harp, harbor and gray seal ... - university of maine
TRANSCRIPT
The University of Maine The University of Maine
DigitalCommons@UMaine DigitalCommons@UMaine
Electronic Theses and Dissertations Fogler Library
Summer 8-22-2020
Harp, Harbor and Gray Seal Strandings in the Gulf of Maine: A Harp, Harbor and Gray Seal Strandings in the Gulf of Maine: A
Retrospective Socio-Ecological Analysis Retrospective Socio-Ecological Analysis
Holland Haverkamp University of Maine, [email protected]
Follow this and additional works at: https://digitalcommons.library.umaine.edu/etd
Recommended Citation Recommended Citation Haverkamp, Holland, "Harp, Harbor and Gray Seal Strandings in the Gulf of Maine: A Retrospective Socio-Ecological Analysis" (2020). Electronic Theses and Dissertations. 3310. https://digitalcommons.library.umaine.edu/etd/3310
This Open-Access Thesis is brought to you for free and open access by DigitalCommons@UMaine. It has been accepted for inclusion in Electronic Theses and Dissertations by an authorized administrator of DigitalCommons@UMaine. For more information, please contact [email protected].
HARP, HARBOR AND GRAY SEAL STRANDINGS IN THE GULF OF MAINE:
A RETROSPECTIVE SOCIO-ECOLOGICAL ANALYSIS
By
Holland Haverkamp
B.A. Brooks Institute of Photography, 2005
A THESIS
Submitted in Partial Fulfillment of the
Requirements for the Degree of
Master of Science
(in Ecology and Environmental Sciences)
The Graduate School
The University of Maine
August 2020
Advisory Committee:
Kristina Cammen, Assistant Professor of Marine Sciences, Advisor
Damian Brady, Associate Professor of Marine Sciences
Sean Todd, Professor of Marine Sciences, College of the Atlantic
© 2020 Holland Haverkamp
All Rights Reserved
HARP, HARBOR AND GRAY SEAL STRANDINGS IN THE GULF OF MAINE:
A RETROSPECTIVE SOCIO-ECOLOGICAL ANALYSIS
By Holland Haverkamp
Thesis Advisor: Dr. Kristina Cammen
An Abstract of the Thesis Presented in Partial Fulfillment of the Requirements for the
Master of Science (in Ecology and Environmental Sciences)
August 2020
Over the past several decades, the Gulf of Maine (GOM) has experienced significant socio-ecological
change. Extreme climatic variation increases in human population, and visitation of coastal areas have
significantly impacted coastal ocean health and redefined multispecies ecologies. While pinniped
populations in the Northeast United States have generally grown following federal protection, they have
also experienced multiple mortality events over the past two decades. Long-term datasets from marine
mammal stranding networks represent a valuable resource for investigating trends in marine mammal
health during this period of change. Here, I evaluated potential drivers of marine mammal strandings
using data collected from stranded harbor (Phoca vitulina), harp (Pagophilus groenlandicus) and gray
(Halichoerus grypus) seals from 2002 to 2017 in Massachusetts, New Hampshire and Maine. I tested for
spatio-temporal correlations between stranding density and potential social (e.g., population density)
and environmental (e.g., sea surface temperature, North Atlantic Oscillation, snowfall and sea ice
extent) factors. Our models reveal significant effects of location and human population density on
stranding rates across species—signifying that, even after correcting for reporting effort, pinnipeds are
more likely to strand near more densely populated human epicenters in the GOM—as well as species-
specific relationships with some environmental factors. These analyses increase our understanding of
the circumstances that lead pinnipeds to strand in the Gulf of Maine and provide context within which
these species may serve as sentinels of coastal ocean health.
i
TABLE OF CONTENTS
LIST OF TABLES………………………………………………………………………………………………………………………….iii
LIST OF FIGURES………………………………………………………………………………………………………….…….……..iv
Chapter
1. INTRODUCTION……………………………………………………………………………………………….……………..1
Study area and species…………………………………………………………………………………………………..3
Harbor seals…………………………………………………………………………………………………………………..5
Gray seals………………………………………………………………………….……………………………………………6
Harp seals………………………………………………………………………………………………………………………8
Stranding data…………………………………………………………………………………………………………….…9
2. METHODS……………………………………………………………………………………………………..……….….…10
Study design………………………………………………………………………………………………………….……..11
Explanatory variables……………………………………………………………………………………………..…….13
Model description……………………………………………………………………………………………………..…17
3. RESULTS……………………………………………………………………………………………………………….………19
4. DISCUSSION………………………………………………………………………………………………………………….28
A tale of two species: seals and humans……………………….…………………………………………..…28
Environmental variables………………………………………….……………………………………………………31
Stranding data: A cautionary tale…………………………………………………………………………………33
5. REFERENCES………………………………………………………………………………………….…………….……….36
6. APPENDICES…………………………………………………………………………………………………………………44
ii
Appendix A: Stranding response organizations…………………………………………………………….44
7. BIBLIOGRAPHY OF THE AUTHOR…………………………………………………………..………………………45
iii
LIST OF TABLES
Table 2.1. Explanatory variables……………………………………………………………………………………………14
Table 3.1. Number, sex, and age class of harbor, harp and gray seal strandings.…….……………19
Table 3.2. Generalized Additive Mixed Model statistics for all models (harbor seal pups,
harbor seal adults, gray seals, harp seal yearlings and harp seal all age classes [AAC])…………….21
Table 3.3. R2 (adjusted) and deviance explained for 5 species/age classes of observed
pinniped strandings in the Gulf of Maine from 2002-2017……………………………….………………………24
iv
LIST OF FIGURES
Figure 1. Map of the Gulf of Maine, including border between US and Canada ………..…………5
Figure 2. Maps portraying stranding density of five pinniped species/age classes.………….…13
Figure 3. Annual strandings of 3 species of seals in the Gulf of Maine from 2002 to 2017.…20
Figure 4. Density maps and smoother estimates of pinniped strandings and covariates.…..26
1
INTRODUCTION
Pinniped abundance and distribution are influenced by a variety of human-related and
environmental factors; however, accurately describing these trends can be difficult, costly and
time consuming as these species spend much of their time at sea (Meager & Sumpton, 2016).
Long-term data collected by marine mammal stranding response programs can be leveraged to
help address these knowledge gaps. Stranding data can offer demographic (Mannocci et al.,
2012) and species diversity information (Pyenson, 2011) that is often lacking in landscape
ecology studies1, thereby enriching our understanding of both species abundance and
distribution as they vary over time and space. Spatio-temporal patterns of strandings can also
provide valuable insight into the varied and interacting factors that influence when, where and
why marine mammals strand.
This type of information can be valuable to agencies involved in marine mammal
management and conservation, as a means to anticipate shifts in marine mammal populations
(Laidre et al., 2015), whether driven by human causes, environmental change, or a combination
of the two. Climate change related range shifts have been observed in many marine mammal
populations (Clarke et al., 2013; Hamilton, Lydersen, Ims, & Kovacs, 2015; Ijsseldijk et al., 2018),
and it is predicted that as the climate progressively changes, these influences will be more
widespread. Marine mammals are widely recognized as indicator species for ocean—and
therefore global—health (Simeone, Gulland, Norris, & Rowles, 2015). They are considered
sentinel organisms because they have long life spans, feed at high trophic levels, have extensive
1 Studies in landscape ecology focus on the patterns and interactions between ecosystems within a region of interest, as opposed to individual species or ecological processes.
2
fat stores and they accumulate anthropogenic toxins (Reddy, Dierauf, & Gulland, 2001). They
are also conspicuous (generally), and hold charismatic value to humans; therefore, they are
more likely to be observed (Bossart, 2011). As climate-induced changes to environmental
health continue, the potentially negative effects on marine mammals, such as epizootic disease
outbreaks, can serve as bellwethers for not only ocean health, but also human health (Bossart,
2011).
Previous studies have found that stranding densities can be predicted in part by
environmental and ecological factors. Studies of stranded pinnipeds, as well as cetaceans, have
found correlations of stranding density with oceanic conditions, such as sea surface
temperature (Ijsseldijk et al., 2018; Macleod et al., 2005), sea ice extent (Johnston, Bowers,
Friedlaender, & Lavigne, 2012; Soulen, Cammen, Schultz, & Johnston, 2013), El Niño and La
Niña (Colegrove, Greig, & Gulland, 2005; Hanni, Long, Jones, Pyle, & Morgan, 1997), and the
North Atlantic Oscillation (Pierce, Santos, Smeenk, Saveliev, & Zuur, 2007; Truchon et al., 2013).
Prado et al. (2016) found that strandings along the east coast of South America were strongly
correlated with seasonality, and they theorized this was an indirect result of fishing effort
impacting cetaceans and post-reproductive dispersal among otariids. However, numerous
studies have also found that variation in stranding frequency and distributions can at least
partially be explained by reporting effort, as this can vary between years and response agencies
(Gulland & Hall, 2007; Papastavrou, Leaper, & Lavigne, 2017; Savenkoff et al., 2007).
Although several studies have used strandings data to analyze abundance and distribution
of seals in the US Gulf of Maine (Harris & Gupta, 2006; McAlpine, Donald F., Stevick, Peter T.,
Murison, 1999; Soulen et al., 2013; Stevick & Fernald, 1998), few have looked at the
3
interconnectedness between anthropogenic and environmental factors influencing when and
where seals strand. Here, I use generalized additive mixed models (GAMMs) to analyze the
harbor (Phoca vitulina), harp (Phoca groenlandica) and gray seal (Halichoerus grypus) stranding
record in the Gulf of Maine from 2002-2017 to better understand how anthropogenic and
environmental factors, specifically human population, sea surface temperature, the North
Atlantic Oscillation, snowfall and sea ice extent in the Gulf of St. Lawrence, influence seal
stranding patterns. Our findings, that pinniped strandings in the Northwest Atlantic are
observed most frequently at human population epicenters, independent of reporting effect,
and that sea surface temperature and the North Atlantic Oscillation may have some predictive
power, provide insights that are relevant to marine mammal policy.
Study area and species
Bordered by Cape Cod, Massachusetts to the south and Nova Scotia, Canada to the
north, the Gulf of Maine (GOM) is a biogeographically distinct province (Byrd et al., 2014).
Topographical features, temperature gradients, and ocean currents that limit recruitment and
affect mortality define marine biogeographic boundaries that are known to have long-term
influences on phylogeography and species diversity within their environments (Wares, Gaines,
& Cunningham, 2001). These environmental discontinuities can have long term impacts on the
ecological landscape. In the Gulf of Maine, Georges Bank, the Scotian Shelf and the Eastern
Maine Coastal Current create environments that are biologically rich, creating what have been,
historically, productive fishing grounds for marine mammals and humans alike.
Concomitant to the long-term effects of these biogeographic features are the relatively
recent—but potentially highly impactful—effects of socio-ecological stressors, such as
4
anthropogenic climate change, which also influence the ecology in the Gulf of Maine. Sea
surface temperature (SST) in the Gulf of Maine is increasing at one of the fastest rates globally
(Pershing et al., 2016), and alteration of SST phenology has extended the summer season by as
much as two days per year over the last thirty years (Thomas et al., 2017). Extent of sea ice in
the Gulf of St. Lawrence has decreased significantly over the last several decades (Ruest et al.,
2015), directly affecting the ecological landscape in the Gulf of Maine through shifts in the
timing of seasonal migrations. The North Atlantic Oscillation (NAO), which has been shown as a
driver of a rapidly changing climate (Delworth et al., 2016), has undergone marked variability
over the last 4 decades (Li, Sun, & Jin, 2013). Simultaneously, tourism in the region has
continuously increased, particularly in the summer months, bringing waves of people to already
contested coastal landscapes, where a legacy of fisheries and other maritime industries are in a
state of flux.
This region, which comprises over 4,000 kilometers of coastline, including inlets and
islands, encompasses all breeding habitats of harbor and gray seals in US Atlantic waters (Figure
1). The southeastern half of this region is made up of sandy coastline and substantial human
development, whereas the northeastern half consists of mostly rocky shores and is
considerably more rural. Dense human population centers include Boston, Massachusetts and
Portland, Maine. Active maritime industries and tourism dominate much of the coastal
landscape, as well as the nearshore waters. Both fisheries and tourism experience strong
seasonal trends. For example, Acadia National Park (in Downeast Maine) brings in over 2.5
million visitors per year, predominantly in the summer months. Cape Cod, Massachusetts
experiences similar trends. In addition to impacting the potential levels of reporting by the
5
public, these strong fluctuations in the phenology of human activity in these environments
directly influence the local ecology, including the local pinniped populations.
Harbor seals
Harbor seals, the most abundant pinniped species in the GOM, inhabit the coastal
waters of Eastern Canada and Maine year-round, but their numbers generally increase from
spring through autumn when thousands migrate to the Northeastern US (Katona, Richardson, &
Rough, 1993). It is during this time, from mid-April to mid-June, when adult females seek out
protected areas to give birth to their pups. As autumn approaches, the seals migrate south to
the Cape Cod region, with hundreds to thousands going as far as North Carolina. This migration
then reverses in spring, and the harbor seals come back to Maine, New Hampshire and Eastern
Canada to spend the summer. During the late 1800’s and well into the 1900’s, harbor—as well
as gray—seal bounties caused the populations to be severely depleted, and even extirpated in
6
several localities. Lelli, Harris and Aboueissa (2009) estimate that roughly 40,000 seal bounties
were collected during the late 19th and early 20th centuries. It was not until after these bounties
were lifted, and the US Marine Mammal Protection Act (MMPA) was passed, that these
populations rebounded (Roman et al., 2013).
arbor seal abundance in Maine increased by 5.5% year-1 after the passage of the MMPA,
with the majority of that increase being pups, which increased from 6.4% of the population in
1981 to 24.4% of the population in 2001 (Gilbert, Waring, Wynne, & Guldager, 2005). As
abundance has increased, so have the number of ledges used during pupping season,
signifying an expansion of distribution during the summer months. More recent
population estimates suggest a leveling off or potential reversal of population growth trends
from the prior decades. Estimates from an aerial survey conducted in 2012 suggested a
decrease in seals from 99,340 in 2001 to 75,834 in 2012 (Waring, DiGiovanni Jr., Josephson,
Wood, & Gilbert, 2015). However, variation in methods between the 2001 and 2012 surveys
and the lack of more recent data (estimates from an aerial survey conducted in 2018 are
pending) have led to uncertainty around the current harbor seal population status.
Gray seals
Gray seals have a more northern distribution than that of the harbor seals, occurring
from Nantucket Sound, Massachusetts, as far north as northern Labrador, Canada (Katona et
al., 1993). The western Atlantic stock breeds in eastern Canada and the northeastern United
States from mid-December to early February. For much of the 20th century, gray seals were
nearly extirpated from US waters, largely due to a lack of protection and aggressive bounties
(Wood, Murray, Josephson, & Gilbert, 2020). Similarly, in Eastern Canada, gray seal populations
7
declined to fewer than 10,000 beginning in the late 1800’s and persisting until the 1960’s
(Lavigueur & Hammill, 1993). More recently, since the cessation of bounties and
implementation of federal protection in US waters, gray seal populations across the Northwest
Atlantic have experienced population growth. The population in Eastern Canada reached an
estimated size of nearly half a million individuals in 2011, and gray seal populations have grown
substantially in abundance in the Gulf of Maine (Hayes, Josephson, Maze-Foley, & Rosel, 2017).
In Maine, haul out sites which were once dominated by harbor seals are now shared with gray
seals (Gilbert et al., 2005). Prior to 1993, no gray seals were observed in aerial surveys
conducted during harbor seal pupping season, but nearly 2,000 were observed in a 2001
survey.
This shift in species composition has been even more dramatic on Sable Island, Canada,
150 miles off the coast of Nova Scotia. Here, gray seals populations have increased
dramatically, and harbor seals have declined to become virtually absent from the colony. Sharks
represent a source of natural mortality in this region, specifically on the smaller harbor seals;
and the rate of shark-induced mortality increased concomitantly with the decrease in harbor
seal abundance during the 1990’s (Lucas & Stobo, 2000). However, shark induced-mortality
alone is not enough to explain the decrease in harbor seals in Eastern Canada. It is feasible that
interspecific competition with gray seals (Hall & Kershaw, 2012; Johnston et al., 2015), which
have overlapping diets, could have caused the harbor seals to decline (Pace et al., 2019; Bowen
& McMillan, 2003). There is evidence that dispersal of gray seals from Sable Island has played a
role in the reestablishment of US pupping sites (Pace et al., 2019), and similar instances of
harbor seals being displaced by gray seals at beaches and ledges have been observed in the
8
Northeast US (Pace et al., 2019). However, the increasing trend of gray seals in Sable Island, as
well as that in Cape Cod, Massachusetts, has slowed compared to a decade ago (M. O. Hammill,
Heyer, Bowen, & Lang, 2017).
Harp seals
The northwest Atlantic harp seal has a complex migration and reproductive cycle.
During winter, they breed on pack ice in the Gulf of St. Lawrence and off Labrador, in Canada.
As the ice retreats in late spring, the seals advance northwards, arriving in Baffin Island and
southern Greenland (Katona et al., 1993). After summer, harp seals then head south again,
ahead of the advancing ice. Although it is beyond the range of the larger colonies, individual
seals do stray into the Gulf of Maine, and occasionally as far south as Virginia. This population
has been commercially harvested since the 1700’s (Sergeant, 1991), and concerns over its
future was one of the factors that contributed to the adoption of the MMPA (Hammill et al.,
2015). The MMPA, combined with a ban on the import of pelts and hunting quotas in Canada
(Katona et al., 1993), as well as a shift in policy and attitudes in Canada, caused their population
to rise from a low of 1.1 million in the early 1970’s to over 7 million in the last decade (Mike O.
Hammill et al., 2015). Before 1994, there were no confirmed harp seal sightings in the Gulf of
Maine; however, since then, sightings have consistently increased, possibly as a result of range
expansion or changing oceanographic conditions (Stevick & Fernald, 1998). It has been shown
that harp seals, particularly yearlings, strand more frequently during years of decreased ice
cover (Soulen et al., 2013). With sea ice generally breaking up earlier in the year as the global
climate warms, pagophilic seals will increasingly spend more time at sea, and it is probable that
they will be more frequent visitors to the Gulf of Maine.
9
Stranding data
In the United States, a national marine mammal stranding network was formed in 1992 as
part of the reauthorization of the US Marine Mammal Protection Act (MMPA). This Act broadly
aims to maintain marine mammal stocks as functional elements in the ecosystem. Towards this
aim, the Marine Mammal Health and Stranding Response Program was created to collect and
disseminate data, correlate the health of marine mammals with environmental parameters,
and coordinate an effective response to unusual mortality events2 (Hofman, 1987; Simeone et
al., 2015). In application, a major responsibility of this program is to respond to stranded
marine mammals. Under section 401(3) of the US MMPA, marine mammals are considered
stranded either when they are dead, or when they are alive and: a) unable to return to the
water, b) in apparent need of medical assistance, and/or c) unable to return to their habitat.
This policy, by prohibiting any incidental takes (“takes” are defined as: to harass, hunt, capture,
or kill, or attempt to harass, hunt, capture, or kill any marine mammal) of marine mammals, is
among the most sweeping environmental policies in modern American history, and resulted in
significant increases in many marine mammal populations—including harbor, harp and gray
seals (Roman et al., 2013). In this study, I aggregated and analyzed the stranding data of harbor,
harp and gray seals in Maine, Massachusetts and New Hampshire from 2002-2017, to better
understand a) their abundance and distribution over the study period and b) what, if any,
environmental and social variables effected where and when strandings were observed.
2 An Unusual Mortality Event (UME) is defined under the Marine Mammal Protection Act” as a stranding event that is unexpected, involves a significant die-off of any marine mammal population, and demands immediate response.”
10
METHODS
Stranding data for this study were extracted by request from the Marine Mammal
Health and Stranding Response Program’s National Stranding Database which includes
contributions from 11 organizations in Maine, New Hampshire and Massachusetts. Contributing
organizations included (from north to south) the College of the Atlantic’s Allied Whale, National
Marine Fisheries Service, Maine Department of Marine Resources, Marine Mammals of Maine,
University of New England Marine Animal Rehabilitation Center, Marine Animal Lifeline,
Seacoast Science Center, New England Aquarium, National Aquarium in Baltimore, International
Fund for Animal Welfare, Riverhead Foundation, and the National Aquarium in Baltimore.
Contact details for these organizations can be found in Appendix A.
The data that these stranding networks collect varies in both complexity and detail, the
most basic being “Level-A Data”, a benchmark that is minimally collected for all stranding
events. Level-A data include date, species, morphology, health/condition, physical evidence of
‘human interaction’ and location of stranding. These data detail, to whatever extent possible,
the circumstances surrounding the marine mammal stranding. In this study, we analyzed 9,165
records of Level-A data from harbor, harp and gray seal strandings that occurred from 2002 to
2017. Although previous studies have utilized this type of data, this is, to my knowledge, the
most extensive analysis of marine mammal stranding data in the Gulf of Maine region to date.
I conducted a hierarchical quality assessment/quality control analysis on the location
information associated with the records, as this information was critical to our spatial analysis.
Location information for strandings is recorded by town and county name, as well as with
latitude and longitude coordinates. These coordinates were first used to plot all points on a
11
map using ArcGIS or Google Earth. This allowed for a visual inspection of outliers, such as points
that were too far from the coast or located outside of the Gulf of Maine. The outliers (n = 121;
1.4% of all strandings) were removed from our analysis. After visual analysis, I then further
inspected a random 10% of the records from each species to ensure the coordinates matched
the locality information provided. Of the records randomly sampled, fewer than 7% had errors
in latitude and longitude coordinates.
When a stranding event is entered into the National Database, an associated confidence
code: low, medium, high or unconfirmed, is chosen based on how confident the reporter is in
the information provided. Observations with unconfirmed confidence codes (n = 621) were not
included in this analysis. Furthermore, any stranding listed with a body condition of
‘mummified’ (n = 170) was not included, because the temporal scale of the analysis might not
accurately reflect the time of death of that seal given its advanced level of decomposition.
Finally, a small sample of harp seal strandings from Massachusetts (n = 33) were not included in
the analysis because they were sourced as part of another study reported by a scientist carrying
out a study on Nantucket Island, rather than by reports to the stranding networks listed above.
After these steps, our final dataset consisted of 8,220 observations.
Study Design
The data were aggregated into 5 separate datasets for analysis: harbor seal adults,
harbor seal pups, harp seal yearlings, all age classes (AAC) of harp seals and all gray seals. These
distinctions were made to better reflect the natural history of each species and age class, with
an aim at understanding how and when they strand, as well as how the circumstances of their
stranding are affected by social and environmental factors. Harp seals, for example, have very
12
different seasonal and temporal migratory patterns than harbor seals, and therefore utilize the
Gulf of Maine in different seasons and in different areas than harbor seals do. Additionally,
these distinctions in datasets were made based on available sample sizes. Gray seals, for
example, could not be parsed into separate datasets based on age class because there were too
few strandings.
My study area was parsed into 0.2° grids (Figure 2). Although a variety of grid sizes were
initially explored (0.05°, 0.1°, 0.4°), this size was ultimately used based on knowledge of the
daily behavior of the pinniped species focused on in this study, and the relative size of the
inlets, bays and islands along the coastal region in our study area. All analyses were completed
at a seasonal time scale where Winter included December, January and February; Spring
included March, April and May; Summer included June, July and August; and finally, Fall
included September, October and November. From 2002 to 2017 in total, our analysis included
64 seasons for which a seal stranding could be observed in any particular grid box. Grid boxes
were only included in the models if there was at least one stranding of that particular
species/age class in any given season over the 16-year time period; therefore, the number and
location of boxes differ between models. For example, when modelling gray seals, if a certain
grid box had 2 records of strandings in Spring 2004, but no other strandings in that grid box
over the 16-year study period, then it would receive a 2 for that box in Spring 2004, and 63 0’s
for the rest of the seasons in that box. Alternatively, if a grid box had no recorded strandings
over the 16-year period it was excluded from the model altogether.
13
Figure 2. Maps portraying stranding density of five pinniped species/age classes. Study region is in the Gulf of Maine from 2002-2017. Grid size is 0.2°.
Explanatory Variables
Based on a combination of ecological relevance and data availability, covariate
exploration yielded inclusion of the following in my analyses: human population density, NAO,
SST, previous season SST, snowfall and sea ice extent (Table 1). Latitude and longitude were
also included as covariates, and year as a random effect. Variance inflation factors were
calculated for all covariates and indicated that correlations between covariates were not a
cause of concern, with the exception of longitude and human population, which had a
threshold greater than 3 (Zuur, Leno & Elphick, 2010). For this reason, longitude was not
included in the models and, instead, human population and latitude were included as an
interacting term.
14
Table 2.1. Explanatory variables. Environmental and social variables utilized in generalized additive mixed models, their source, raw geographic range and raw temporal scale.
Variable Source Scale and Resolution (Raw Data)
Geographic Temporal
Environmental
Sea surface temperature Satellite Oceanography Data Laboratory, University of Maine
1.1 kilometer Daily
Sea Ice Cover NASA Sea Ice Concentrations - Nimbus-7 SMMR and DMSP SSM/I-SSMIS Passive Microwave Data algorithms
Gulf of St Lawrence Monthly
NAO Index NOAA Climate Prediction Center
North Atlantic Monthly
Snowfall Northeast Regional Climate Center, Cornell University
Variable locations Daily
Social
Human population density US Census Bureau Coastal towns of ME, NH, MA Annual
Human population data were procured from the US Census Department, and
aggregated by year and by town for all towns that contained at least one stranding over the
time series. After correcting town names that were duplicates of each other in the stranding
database, but with minor disparities (e.g., Addison vs. Addison Town), there were 253 towns in
Maine, 155 in Massachusetts, and 49 in New Hampshire, for a cumulative total of 457 towns in
our dataset. Final values used in analysis were the sum of census counts for all towns in a given
year in a particular grid box. Where values were missing because a grid box did not contain any
towns, an average of nearest neighbor values was used. Nearest neighbors in this case refers to
any grid box surrounding the grid box with a missing value, or approximately a circle with a
radius of 29km. Population values were converted to a log scale for analyses, to correct for
skewness created by large values, such as in Boston, Massachusetts or Portland, Maine.
15
I utilized NAO index data from the National Oceanic and Atmospheric Administration
(NOAA), Climate Prediction Center (“Daily North Atlantic Oscillation Index,” 2002). The NAO
index is a measure of the sea-level pressure difference in the North Atlantic Ocean between the
Subtropical High and the Subpolar Low. A negative NAO pressure value, which represents
relatively small differences between these two pressure gradients, is typically conducive of
colder, wetter winters in the Northeast US. This index serves as a proxy for climatic variability
over the entirety of the North Atlantic Ocean, and several studies have found significant
correlations between it and marine mammal strandings (Evans et al., 2005; Truchon et al.,
2013). Furthermore, this cyclical climatic variation has been linked with recruitment of multiple
pagophilic seal species (Ferguson, Stirling, & McLoughlin, 2005; Friedlaender, Johnston, Fink, &
Lavigne, 2006), positioning it as an important explanatory variable for this study. The
standardized anomalies are calculated and collected by NOAA Fisheries, and therefore no
further manipulation of the raw data were required for our analysis other than to convert the
monthly values into seasonal averages.
NOAA satellite SST data were received, processed and provided by Dr. A. Thomas,
Satellite Oceanography Data Lab, University of Maine. Observations were made daily at a
spatial scale of 1.1km, and converted into seasonal anomalies to coincide with our study
parameters. Nearest neighbors (average of all data points contiguous to the missing value) and
nearest-neighbors’ neighbors (average of data points abutting nearest neighbors) were used to
fill in missing values, when possible (e.g., missing due to cloud cover). Grid boxes for which SST
could not be imputed in this fashion (~1% of grid boxes for the harbor seal pup and adult
models) were excluded from the analysis so that sample sizes were equal across all models and
16
AIC values were comparable. Using a cross correlation function, I identified that the strongest
correlation between SST and stranding density in our dataset occurred at a 4-month lag; that is,
the probability of a stranding being observed as a function of SST was most affected by values
four months before that stranding. For that reason, SST for the season before the observed
stranding (“prev SST”) was also included in our models. SST has been correlated with frequency
of marine mammal stranding in all parts of the globe and across most marine mammal taxa
(Forcada, Trathan, Reid, & Murphy, 2005; Ijsseldijk et al., 2018; Macleod et al., 2005; Truchon et
al., 2013).
It has been shown that pagophilic seals occasionally consume snow, presumably for the
sake of hydration (Schots, Bue, & Nordøy, 2017), when other forms of freshwater are scarce—
potentially situating snow as a limiting resource during harp seal migration. Snowfall data were
collected by the Northeast Regional Climate Center of Cornell University. From raw daily
snowfall values, I calculated cumulative monthly values in each grid box. In the event a grid box
did not have a snowfall value, nearest neighbors and nearest-neighbors’ neighbors were used,
as described above. These monthly cumulative totals of snowfall were then converted into
monthly anomalies. The three-monthly anomalies in a given season were then averaged to
create one seasonal value per grid box.
Hammill et al. (2015) found that poor sea ice conditions result in increased harp seal
pup mortality, particularly if a threshold level of 60% decline in sea ice cover is met. Sea ice
coverage data used in this study were produced by the US National Sea Ice Data Center in
Boulder, Colorado. Given the seasonality of harp seal breeding, pupping and southern
migration, only values during the winter and spring were utilized. The sea ice coverage values
17
were derived from the Defense Meteorological Satellite Program’s Special Sensor Microwave
Imagers (satellites F8, F11, and F13) for 2002 through 2007 and Special Sensor Microwave
Imager Sounder (satellites F16, F17 and F18) for 2008 through 2017. Monthly mean values were
used to create seasonal averages, resulting in a single value for ‘winter’ and a single value for
‘spring’ which were used in the harp seal models, regardless of which grid box a stranding was
observed in.
Model Description
Generalized Additive Mixed Models (GAMMs) were used to analyze the relationship
between the frequency of strandings in a grid box (with no observations being a ‘0’, a single
stranding in one grid box in one season being a ‘1’, and so on) in a season and the explanatory
variables using a tweedie distribution model. A tweedie model was utilized due to its ability to
handle a substantial number of 0’s in the data (Tweedie, 1984), as is the case in this study since
observed strandings can be scarce, particularly in more rural areas or outside of the seals’
migratory seasons. GAMMs are a useful tool here because they combine the use of linear mixed
models, which incorporate random effects, and generalized linear models, which can handle
non-normal data (Bolker et al., 2009). Additionally, this function allows for cross validation,
which automatically determines the optimal amount of smoothing, capturing important
patterns in the data (Zuur et al., 2009). The full GAMM, evaluated independently for each of
five models—harbor seal adults, harbor seal pups, harp seal yearlings, harp seal AAC, and gray
seals—included the variables latitude, season, human population, human population:latitude,
SST for the current and previous seasons, NAO, and a random effect for year. To account for the
time they spend in the GOM (either due to migration patterns or pupping season), harp seal
18
models (for yearling and all age classes) and harbor seal pup models were limited to two
seasons—winter and spring for harp seals, and spring and summer for harbor seal pups. The
harp seal models (yearlings and AAC) also incorporated the variables snowfall and sea ice
extent. Human population and latitude were included in all models as control variables. Human
population in particular was used as a correction term for sighting probability (i.e., observation
effort). All modeling was completed using the ‘mgcv’ package in R Studio version 1.2.5 (R
Development Core Team 3.0.1., 2013).
‘Year’ was treated as a random effect to account for the effects of episodic or sporadic
events that could not be included in our model, such as unusual mortality events (UMEs). 2006,
for instance, had nearly three times greater strandings than the average of all years over the
study period. During this time, NOAA Fisheries had declared an UME for pinnipeds between
Virginia and Maine; in total, an estimated 800 pinnipeds were identified as part of this UME. A
similar UME occurred in 2011, affecting 784 pinnipeds in Maine, New Hampshire and
Massachusetts. Infectious disease was determined to be the cause in both of these cases.
Modelling within each of the five datasets was done in a stepwise fashion, beginning
with a base model (human population:latitude, human population, latitude and year), and then
incrementally adding the remaining explanatory variables one at a time and cumulatively until
all combinations had been explored. “Deviance explained” (analogous to variance in a linear
regression), adjusted R2, and Akaike Information Criterion (AIC) scores were calculated.
Smoother estimates for the selected covariates were plotted. When the slopes were positive,
the covariates were related positively to the dependent variables, suggesting that an increase in
the explanatory variable correlates with an increase in stranding density.
19
RESULTS
From 2002 to 2017, local marine mammal stranding response networks identified and
recorded 9,165 stranded harbor, harp and gray seals in the Gulf of Maine between
Massachusetts and Maine. Of these 9,165 records, 8,220 were considered viable for this study
following the quality control/quality assessment procedures described above. The majority
(69.0%) of stranded pinnipeds in our study area were harbor seals (Table 2). The most
commonly stranded age class per species were pups (66.0%) for harbor seals, yearlings (69.8%)
for harp seals, and adults (31.1%) for gray seals. Males stranded more frequently than females
in all species, particularly with the harp seals, where 47.9% were males, 27.4% were females,
and 24.8% could not be identified.
Table 3.1. Number, sex, and age class of harbor, harp and gray seal strandings. Study area is Maine, New Hampshire and Massachusetts from 2002 to 2017 (N=8,220).
Total strandings Sex (%/Species) Age Class (%/Species)
Species (n) (%) Male Female Unk. sex Pup Yearling Subadult Adult Unk. age
Harbor seal 5,666 69.0 32.2 30.5 38.2 66.0 9.4 4.7 15.1 4.8
Harp seal 1,277 15.5 47.9 27.4 24.8 1.2 69.8 10.8 8.5 9.7
Gray seal 1,277 15.5 41.6 32.3 26.2 24.1 17.1 20.8 31.1 9.9
The frequency of gray seal strandings increased significantly over the study period, from 17 in
2002 to 168 in 2017, whereas the frequency of harp seal strandings decreased significantly,
from 89 in 2002 to 36 in 2017 (Figure 3). Harbor seal stranding frequency was relatively flat
over the 16-year period, with the exception of in 2004-2006 and 2011 when a
20
disproportionately high amount stranded due to UME’s, which were declared in 2—6 and 2011.
Harp seals also saw a spike in strandings around that time, in 2004, and saw a general decline in
stranding frequency over the stranding period.
Figure 3. Annual strandings of 3 species of seals in the Gulf of Maine from 2002 to 2017. Dashed lines represent the linear trend for each species.
Final models explained 29.4% to 47.3% of the total deviance in stranding density, with
gray seal models explaining the least and harp seal AAC models explaining the most (Table 3).
The majority of this explained deviance could be attributed to the four parameters included in
the base model for all species and age classes examined here. Total deviance explained in base
models, which include human population, latitude, human population:latitude, and year,
ranged from a low of 29.4% in the gray seal model to a high of 45.8% in the harp seal AAC
model. Year, and the interaction between human population and latitude, were statistically
21
significant predictor variables in all models. When modeled with the random effect year alone,
deviance explained and adjusted R2 were much lower than the base model, ranging from 2.69%
explained in the harbor seal pup model, to 15.4% in the harp seal yearling model.
Table 3.2. Generalized Additive Mixed Model statistics for all models (harbor seal pups, harbor seal adults, gray seals, harp seal yearlings and harp seal all age classes [AAC]). Models included human population density (pop), latitude (lat), the interaction of human population density and latitude (pop:lat), sea surface temperature (sst), sea surface temperature for the previous season (prev sst), North Atlantic Oscillation (nao), snowfall (snow), and sea ice extent in the Gulf of St. Lawrence (ice). Akaike Information Criterion (AIC) scores are presented as differences from the lowest score within each category. Asterisks denote statistical significance (‘<0.1, *<0.05, **<0.01, ***<0.001). Sample size (n) for each model is the product of the number of grid boxes and number of seasons. Model Adjusted R2 Deviance % Δ AIC
Harbor seal - pup, n = 4464
pop:lat***, pop, lat, year*** 0.178 33.2 269.166
pop:lat***, pop, lat, sst**, year*** 0.299 39.7 2.873
pop:lat***, pop, lat, prev sst**, year*** 0.299 39.7 3.129
pop:lat***, pop, lat, nao**, year*** 0.214 35.0 202.521
pop:lat***, pop ,lat, nao*, sst**, year*** 0.302 39.9 1.242
pop:lat***, pop, lat, nao*, prev sst*, year*** 0.302 39.9 0
Harbor seal - adult, n = 4864
pop:lat***, pop, lat*, year*** 0.140 32.5 3092.914
pop:lat***, pop, lat*, sst**, year*** 0.266 39.7 14.882
pop:lat***, pop, lat', prev sst**, year*** 0.276 39.6 36.574
pop:lat***, pop, lat’, nao***, year*** 0.168 34.2 2240.95
pop:lat***, pop, lat*, nao, sst**, year*** 0.266 39.7 10.47
pop:lat***, pop, lat', nao*, prev sst**, year*** 0.283 39.8 0
Gray seal, n = 4992
pop:lat***, pop, lat, year*** 0.157 29.4 0
pop:lat***, pop, lat, sst*, year*** 0.262 37.6 3715.675
pop:lat***, pop, lat, prev sst**, year*** 0.266 37.6 3733.675
pop:lat***, pop, lat, nao, year*** 0.254 37.3 3592.475
pop:lat***, pop, lat, nao, sst**, year*** 0.260 37.6 3740.135
pop:lat***, pop lat, nao, prev sst**, year*** 0.265 37.6 3740.855
Harp seal - yearling, n = 2304
pop:lat***, pop*, lat*, year*** 0.362 43.9 0
22
pop:lat***, pop*, lat*, sst*, year*** 0.368 44.2 90.998
Table 3.2 continued
pop:lat***, pop, lat, prev sst**, year*** 0.361 43.9 1.966
pop:lat***, pop', lat, nao***, year*** 0.382 45 297.742
pop:lat***, pop', lat*, snow, year*** 0.368 44.2 71.929
pop:lat***, pop*, lat*, ice, year*** 0.368 43.9 15.128
pop:lat***, pop*, lat*, nao***, sst, year*** 0.385 45.2 361.886
pop:lat*** ,pop*, lat*, nao***, sst, ice, year*** 0.385 45.1 361.619
pop:lat***, pop', lat*, nao***, sst, snow, year*** 0.385 45.3 432.527
pop:lat***, pop', lat*, nao*** sst, snow, ice, year*** 0.384 45.3 429.599
pop:lat***, pop', lat*, nao***, snow, ice, year*** 0.38 45.2 377.726
pop:lat***, pop', lat*, snow, ice, year*** 0.367 44.1 71.798
pop:lat***, pop', lat*, sst*, snow, ice, year*** 0.372 44.4 146.746
pop:lat***, pop', lat*, nao***, snow, ice, year*** 0.38 45.2 377.726
pop:lat***, pop', lat*, prev sst, snow, ice, year*** 0.366 44.2 81.209
pop:lat***, pop', lat*, nao***, prev sst, snow, ice, year*** 0.38 45.2 380.506
Harp seal AAC, n = 2464
pop:lat***, pop, lat**, year*** 0.405 45.8 0
pop:lat***, pop, lat**, sst**, year*** 0.412 46.1 105.721
pop:lat***, pop, lat, prev sst, year*** 0.403 45.9 5.894
pop:lat***. pop, lat, nao***, year*** 0.423 47.1 475.637
pop:lat***, pop, lat, snow, year*** 0.408 46.1 117.457
pop:lat***, pop, lat**, ice, year*** 0.404 45.9 8.4
pop:lat***, pop, lat**, nao***, sst, year*** 0.424 47 448.873
pop:lat***, pop, lat**, snow, ice, year*** 0.406 46 60.538
pop:lat***, pop, lat**, prev, snow, ice, year*** 0.405 46 66.331
pop:lat***, pop, lat**, sst**, snow, ice, year*** 0.413 46.3 169.354
pop:lat***, pop, lat*, nao***, sst, snow, ice, year*** 0.423 47.3 555.619
Although the environmental variables often showed significant impacts on the
probability of observing a stranded seal, their effect size was relatively small (Table 4). The
environmental variables that increased the total deviance explained by the greatest amount
23
when added to the base model were SST and previous SST, which increased deviance by 6.5%,
7.2% and 8.2% in the harbor seal pup, harbor seal adult and gray seal models, respectively.
These, along with NAO in the gray seal model, which increased total deviance explained by
7.9%, were the only environmental variables that were, perhaps, biologically relevant.
However, NAO was not statistically significant in the gray seal models.
In the harbor seal pup model, both SST and previous SST predicted a doubling of
stranding density, from 0.5 to 1.0 stranding per grid box per season, when temperatures
increased from 0°C to 3°C warmer than the seasonal average (Figure 3). By contrast, the density
of harbor seal adult strandings peaked at an SST anomaly of 0°C, and decreased three-fold
(from 0.15 to 0.05 strandings per grid box per season) as the average seasonal SST increased or
decreased by 3°C. When analyzing with SST for the previous season, the trend was similar but
the peak was at 1.5°C, as well as when SST approached -3°C. Gray seals response to SST
appeared minimal; from -3°C to 3°C, stranding density increased from 0.0 strandings to 0.03
strandings—a very small magnitude. With prev SST, stranding density increased from 10
strandings at -3°C to 15 strandings at 0°C, and then decreased again to 5 at 3°C.
Among the harp seal yearling and AAC models, the only environmental variable that
explained more than 0.3% was NAO, at 1.1% and 1.3% respectively. The relationship between
harp seal stranding density and NAO was bimodal: higher stranding densities were found at
index values of -0.6 and 0.6 (Figure 3). Harbor seal pup and adult strandings were not
correlated strongly with NAO; the deviance explained by those parameters was 1.8% and 1.7%,
and the confidence intervals were relatively wide.
24
Table 3.3. R2 (adjusted) and deviance explained for 5 species/age classes of observed pinniped strandings in the Gulf of Maine from 2002-2017. Base model includes human population:latitude, human population, latitude and year as explanatory variables. Additional explanatory variables equate to the base model plus that covariate alone. Deviance explained values in SST, previous SST, NAO, snowfall and sea ice extent columns are in addition to the value in the base model.
Species Base model SST Previous SST
NAO Snowfall Sea ice extent
Dev % Adj. R2 Δ Dev % Adj. R2 Δ Dev % Adj. R2 Δ Dev % Adj. R2 Δ Dev % Adj. R2 Δ Dev % Adj. R2
Harbor seal pups 33.2 .178 6.5 .299 6.5 .299 1.8 .214 na na na na
Harbor seal adults
32.5 .140 7.2 .266 7.1 .276 1.7 .168 na na na na
Gray seals 29.4 .157 8.2 .262 8.2 .266 7.9 .254 na na na na
Harp seal yearling 43.9 .362 0.3 .368 0.0 .361 1.1 .382 0.3 .368 0.0 .368
Harp seal AAC 45.8 .405 0.3 .412 0.1 .403 1.3 .423 0.3 .408 0.1 .404
The model that explained the greatest deviance in seal stranding densities was the harp
seal AAC model that included human population, latitude, and their interaction, year, SST, NAO,
snowfall and sea ice extent in the Gulf of St. Lawrence. However, at 47.3% deviance explained,
this is only 0.2% more than that same model without sea surface temperature, snowfall and sea
ice extent. Based on AIC scores alone, “best” models were as follows:
• Base model plus prev SST and NAO for harbor seal pups (AIC 8897) and adults (AIC 6999)
• Base model for gray seals (AIC 6540), harp seal yearlings (AIC 5624) and harp seal AAC (AIC 4163).
For the harbor seal models, the base model plus prev SST and NAO also explained the
greatest deviance. In the gray seal models however, utilizing either SST, prev SST, NAO, or a
25
combination of them yielded an extra ~8% deviance explained and a ~0.11 increase in the
adjusted R2 value. Using AIC scores to choose the “best” model, despite having a lower effect
size, is reflective of the optimal tradeoffs between bias and variance (Richards, 2005). Thus one
should decide which model(s) is an oversimplification of the system, and which are too
uncertain due to the additional parameters (Burhnam & Anderson, 2002). Importantly,
Burhnam and Anderson (2002) note that this rationale of minimizing bias and variance is a
statistical concept and not necessarily reflective of a biological [ecological] reality.
The highest density of strandings were observed across all models at the latitudes
where human populations were high (Figure 3). The highest density of harbor seal pup and
adult strandings occurred at a latitude of 43.5°, the location of Portland, Maine, when the
population in a grid box was approximately 100,000 people. Gray seals also exhibited a narrow
peak of high density strandings located further to the south at latitude 42°, in Cape Cod,
Massachusetts, where the population in a grid box was about 10,000. Harp seals exhibited a
bimodal distribution of peak stranding density, with a strong peak in the Portland, Maine region
and a somewhat lesser peak in the Massachusetts region. They also exhibited a unique pattern
of stranding density centered at latitude 43.5°, in which density was markedly high as
population increased in a cone-like shape that became more broad and diffuse as population
increased, signifying that at those higher population values latitude is not as strong a factor.
26
Figure 4. Density maps and smoother estimates of pinniped strandings and covariates. Density maps (left) are of the interaction between human population (log scale) and latitude of stranded pinnipeds. Smoother estimates (solid lines) are for the environmental predictors of sea surface temperature, North Atlantic Oscillation, snowfall and sea ice extent as obtained by generalized additive mixed models (GAMMs) for stranded pinnipeds. Each covariate smoother was chosen from the model that included the base model plus that individual covariate only. The approximate 95% confidence envelopes are indicated (gray shading). * in the top right corner of variables signify that they are statistically significant. Hash marks on bottom of plots represent observations with positive residuals, and those on the top are observations with negative residuals.
Snowfall and sea ice extent in the Gulf of St. Lawrence were only utilized in the harp seal
AAC and harp seal yearling models. The harp seal AAC models generally exhibited a linear
increase in expected strandings as sea ice extent increased, whereas the harp seal yearling
27
models were relatively flat (Figure 3). Both had large confidence intervals (CIs), in which 95% of
the density in strandings was expected to occur (Nakagawa & Cuthill, 2007). In the harp seal
yearling and harp seal AAC models, neither sea ice extent nor snowfall showed substantive
predictive power on stranding density.
28
DISCUSSION
A tale of two species: seals and humans
This study utilized harbor, harp and gray seal strandings data to investigate spatial and
temporal occurrence patterns in the Gulf of Maine over a 16-year period. It further identified
potential links between stranding events and both anthropogenic and environmental
conditions using GAMMs. Our results illustrate the influence of the interaction between human
population density and latitude on stranded seal density. In all models, this relationship
explained more than any other available explanatory variable, including SST, NAO, snowfall, and
sea ice extent. Neither population nor latitude alone explained nearly as much variability as
their combined interaction. From this interaction, I can infer that seals are not only stranding
more frequently in specific geographic regions simply because of where they are, but because
of how the landscape is being utilized by humans. I propose here two hypotheses as to why
seals strand, or why stranded seals are more frequently observed, near more densely
populated centers.
First, when more humans are present there is an increased likelihood that a stranded
seal will be observed (reporting effect), simply because there are “more eyes on the beach.”
This theory is consistent with our study findings, considering that observations of stranded seals
were significantly higher in areas surrounding the urban centers of Portland, Maine and Cape
Cod, Massachusetts and significantly lower in more rural areas, specifically in Eastern Maine.
However, to help correct for this observer bias in data analysis, human population density was
also included as an explanatory variable in all models. As a linear correction term, human
population should correct for increased observation as it relates to higher population levels. Yet
29
still, the interacting term of human population and latitude was a significant predictor of seal
strandings. If population alone had the same level of influence on stranding observations, the
density plot in Figure 2 would have been a gradient with density increasing from left to right.
Similarly, if latitude had the same level of influence, the density plots would have a gradient of
more frequent strandings across all population values at those latitudes where strandings were
most frequently observed.
A second hypothesis proposed here on the link between human population, latitude and
observed seal strandings is that human activities are leading to, or at least influencing, when
and where a seal strands. This interaction term signifies that there are more strandings on a per
capita basis in specific areas. That is to say, if you are on the coast in one of the stranding
hotspots, you are more likely to observe a stranded seal than if you go to the coast in an area
where fewer strandings have been observed. This may seem obvious, but it is an important
distinction—that there are not simply more people in more urbanized areas to observe
stranded seals; there are, instead, a greater number of stranded seals to observe. This line of
inquiry is well supported in both the academic literature (Barcenas-De la Cruz, DeRango,
Johnson, & Simeone, 2017; Moore et al., 2013; Truchon, Measures, Brêthes, Albert, & Michaud,
2018) and in the Level-A datasheets created by the stranding response agencies. All Level-A
datasheets include the presence/absence of Human Interaction (HI), and when present, these
data include a HI Report. Evidence of HI was noted in the Level-A forms for 11.3% (n = 834) of
stranded pinniped cases during the study period. Evidence of human interaction is noted only
when the response team can reasonably assert that human activities were involved in the
stranding, such as when interactions are observed or through physical evidence (i.e. fishing
30
gear, vessel wounds). This conservative approach to noting human interaction therefore likely
underestimates the influence of humans on these seal populations, as there is often no
evidence for an observer or professional marine mammal responder to say with certainty
whether a marine mammal’s stranding was human induced. This is further confounded when
multiple factors lead to a seal’s stranding, as is often the case (e.g. entanglement in debris leads
to poor nutrition, etc.).
It is important to note that the influence of human population and latitude on pinniped
strandings in the GOM represents a strong spatial signal in these two coastal regions (Portland,
Maine and Cape Cod, Massachusetts). Although the generalizability of these results has not
been tested, it is likely that similar findings may be discovered in other coastal human
epicenters. The coastal regions of the Northeast US encompass a contested landscape between
humans and non-humans. The built environment at the land-sea interface has altered any
concept of what was once “pristine.” The structure and function of marine ecosystems, as well
as their ability to recover from anthropogenic and environmental perturbations, have been
altered (Sherman, 2000), especially since colonization and industrialization. Recreation,
tourism, resource use and industry have taken humans well beyond the confines of their
terrestrial base and into the Gulf of Maine itself. Marine vessels (Vanderlaan & Taggart, 2007;
Wilson et al., 2017), noise (Halliday, Insley, Hilliard, de Jong, & Pine, 2017; Koschinski et al.,
2003), pollution (Kucklick et al., 1994; Reijnders, 1986; Swart et al., 1994), toxins and debris
(Engler, 2012; Simmonds, 2017), and competition for prey (Matthiopoulos et al., 2008;
Overholtz & Link, 2007; Read, 2008) are all recognized as potential contributors to declining
marine mammal health. These waters, once dominated by marine mammals and other aquatic
31
organisms are now increasingly shared. In this new ecology, multiple species are inextricably
entangled - influencing each other's health and wellbeing, restricting each other’s survival and
livability, and frequently redefining what it is to be resilient.
Environmental variables
Despite often being statistically significant (p < 0.05), many of the environmental
variables used in this study are unlikely to be biologically relevant. A doctrine that statistical
significance—the ability to reject our null hypothesis—has been given undue importance in the
ecological sciences has begun to pervade science (Nakagawa & Cuthill, 2007). Instead, it is far
more important to consider the strength of the relationships as indicated by the R2 coefficients
and the deviance explained (Martínez-Abraín, 2008). These statistical metrics are more
appropriate for the determination of whether or not an explanatory variable is biologically
relevant; and in the case of this study, the R2 coefficients and the deviance explained were low
for most environmental variables across models.
The strength of the anthropogenic factors on expected deviance in seal stranding
density are so strong that they may, in part, be overshadowing any impact that the
environmental variables have. Both sea ice extent in the Gulf of St. Lawrence (Johnston et al.,
2012; Soulen et al., 2013; Truchon et al., 2013) and NAO (Ari S. Friedlaender, Johnston, &
Halpin, 2010; Johnston et al., 2012; Truchon et al., 2013) have been correlated with pinniped
strandings in other studies. At 7.9%, NAO is, perhaps, relevant in predicting gray seal strandings
in our models; however, a very wide CI and higher AIC score (in relation to the other models)
signify this may not, in fact, be biologically relevant. Harp seals require ice for successful
molting, pupping, nursing and resting; thus a reduction in sea ice is potentially deleterious to
32
their general health and reproductive success. Yet, my models failed to find that either NAO or
sea ice extent had any effect on stranding density. However, I would caution against
straightforward thinking and linear causation in this case. Harp seals are adapted to cope with
environmental variability and may be buffered against variations in climate (Friedlaender et al.,
2010). It is also possible that a loss of sea ice has opened up feeding pathways and increased
productivity, both of which could, potentially, benefit seals in the region. Further confounding
the relationship, sea ice melting sooner might induce earlier harp seal migration, allowing them
to migrate farther than they ever have in recorded history. It may be that they are indeed
stranding more frequently as a result of these changing climatic conditions, but the data are
masked to the constraints of our study area. Related to this, it is plausible that the high mobility
inherent in pinnipeds may allow them to escape adverse environmental conditions by rapidly
responding to the effects of climate change or other disturbances (Harwood, 2001) and escape
the adverse impacts of a fragmented landscape (Debinski & Holt, 2000).
Harbor pup, harbor adult and gray seal models all reflected an effect of SST on stranding
density; SST for the previous season had an even better fit within models than the current
season, although only marginally. MacLeod et al. (2005) found that warming waters lead to a
decline in cold water marine mammal species and an increase in warm water species. Although
their study was limited to dolphins and porpoises, this hypothesis would be consistent with this
study, as SST appears to be linked to harbor and gray seal strandings. It is also notable that harp
seal stranding observations have decreased over the study period, in line with increased sea
surface temperatures. Similarly, Ijsseldijk et al. (2018) contribute shifts in white-beaked dolphin
distribution in the North Sea coast at least partially to anthropogenic climate change and its
33
concomitant effects (habitat suitability, prey distribution and prey availability). The effect of
warming waters in the GOM on harbor and gray seal strandings cannot be analyzed in a
vacuum, as these effects are inextricably linked with anthropogenic forcings, namely a changing
climate – a reflection of a human population ruled by a global, capitalist market.
Although marine mammal distributions may be influenced by oceanographic and
environmental variables, such as those utilized here, it is often believed that marine mammals
do not respond to them directly (Palacios, Baumgartner, Laidre, & Gregr, 2014), if at all. Many
factors: prey availability, socializing, site fidelity, interspecies competition, direct removal (i.e.,
sealing), bycatch, etc., all may be indirectly influenced by environmental conditions and
phenomena. Thus, these variables can be difficult to measure and model. Further complicating
things is that, in marine ecosystems, predictor variables measured in the ‘present’ are often the
manifestation of the past (Olson, 2002), or perhaps situated in the present and multiple pasts,
potentially resulting in spatial and temporal mismatch (Grémillet et al., 2008). All of these
interactions will lead to reduced explanatory power.
Stranding data: a cautionary tale
Marine mammal stranding data have the potential to be highly valuable to aid in our
understanding of threats to individuals (e.g., entanglement), populations (e.g., epizootic disease
outbreaks), and ecosystems (e.g., climate changes). Yet, it is important to note that there are
numerous challenges and potential issues with using strandings data for scientific research. The
consistency of data can vary widely over time; it is opportunistic, making it vulnerable to
reporting bias (Harris & Gupta, 2006). The coastline in the Northeastern US is extensive, and
thus stranding networks rely substantially on public reporting and trained volunteers.
34
Additionally, it is not uncommon for stranding networks to change protocols over time,
particularly as staff and volunteers change (Harris, Lelli, & Jakush, 2002), which can also lead to
inconsistency, non-standardized protocols, and spatial or temporal gaps in reporting. “Carcass
drift” can result in a carcass being discovered far away from where the original mortality event
occurred (Peltier et al., 2014), if at all (Williams et al., 2011), creating ambiguity in both time
and location, and sometimes cause of death. Finally, public reporting of animals on the beach
may not be stranded at all, but could simply be resting, pupping or molting animals, leading to
potential over-representation of observed strandings, particularly in populated areas. Despite
these challenges, strandings provide a unique dataset that would otherwise be difficult and
costly to collect. These data, when continuously collected—as is the case with the data used in
this study—achieve high temporal and spatial resolution, yielding an invaluable resource to
better understand the spatio-temporal patterns in marine mammal distribution and behavior,
as well as how marine mammals are influenced by anthropogenic and environmental factors.
As existing and emerging risks to marine mammals from environmental forcing and
anthropogenic activities are realized, conservation and management-driven spatio-temporal
models that account for these factors are increasingly salient. This study indicates that, in the
GOM, proximity to dense, coastal human population centers is the greatest driver in pinniped
stranding density. SST is also biologically relevant in harbor seal pup and adult stranding
patterns, as is SST and NAO for gray seals. Future studies might consider more creative
approaches to both modeling and methodology, including the use of local wisdoms. As highly
migratory species that cross biogeographical and political boundaries, no one stakeholder
group alone can fully address their health. Considered together, scientific and traditional
35
ecological knowledge can bring fresh perspectives. Successful conservation will require
communication across a diversity of stakeholders that directly engage with the species (e.g.,
local and regional governments, indigenous groups, non-governmental groups), as well as
continued engagement by federal governments.
36
REFERENCES
Barcenas-De la Cruz, D., DeRango, E., Johnson, S. P., & Simeone, C. A. (2017). Evidence of anthropogenic trauma in marine mammals stranded along the central California coast, 2003-2015. Marine Mammal Science, 2003–2015.
Bolker, B. M., Brooks, M. E., Clark, C. J., Geange, S. W., Poulsen, J. R., Stevens, M. H., & White, J.
S. (2009). Generalized linear mixed models: a practical guide for ecology and evolution. Trends in Ecology and Evolution, 24(3), 127–135.
Bossart, G.D. (2011). Marine mammals as sentinel species for oceans and human health.
Veterinary Pathology, 48(3), 676–690. Bowen, W.D., McMillan, J., & Mohn, R. (2003). Sustained exponential population growth of grey
seals at Sable Island, Nova Scotia. ICES Journal of Marine Science, 3139(03), 1265e1274. Burhnam, K., & Anderson, D. (2002). Model Selection and Mulit-Model Inference. In Model
Selection and Multi-Model Inference. 2nd Edition. Byrd, B.L., Hohn, A .A., Lovewell, G. N., Altman, K. M., Barco, S. G., Friedlaender, A. S.,Harms,
C.A., McLellan, W. A., Moore, K. T., Rosel, P. E., & Thayer, V. G. (2014). Strandings as indicators of marine mammal biodiversity and human interactions off the coast of North Carolina. Fishery Bulletin, 112(1).
Clark, W. (2010). Principles of landscape ecology. Nature Education Knowledge, 3(10), 34. Clarke, J., Stafford, K., Moore, S. E., Rone, B., Erts, L., & Crance, J. (2013). Subarctic cetaceans in
the southern Chukchi Sea: Evidence of recovery or response to a changing ecosystem. Oceanography, 26(4), 136–149.
Colegrove, K. M., Greig, D. J., & Gulland, F. D. (2005). Causes of Live Strandings of Northern
Elephant Seals (Mirounga angustirostris) and Pacific Harbor Seals (Phoca vitulina) Along the Central California Coast, 1992-2001. Aquatic Mammals, 31(1), 1–10.
Daily North Atlantic Oscillation Index. (2002). Debinski, D. M., & Holt, R. D. (2000). A survey and overview of habitat fragmentation
experiments. Conservation Biology, 14(2), 342–355. Delworth, T. L., Zeng, F., Vecchi, G. A., Yang, X., Zhang, L., & Zhang, R. (2016). The North Atlantic
Oscillation as a driver of rapid climate change in the Northern Hemisphere. Nature Geoscience, 9(7), 509–512.
37
Engler, R. E. (2012). The complex interaction between marine debris and toxic chemicals in the
ocean. Environmental Science and Technology, 46(22), 12302–12315. Evans, K., Thresher, R., Warneke, R. M., Bradshaw, C. A., Pook, M., Thiele, D., & Hindell, M. A.
(2005). Periodic variability in cetacean strandings: links to large-scale climate events. Biology Letters, 1(2), 147–150.
Ferguson, S. H., Stirling, I., & McLoughlin, P. (2005). Climate change and ringed seal (Phoca
hispida) recruitment in western Hudson Bay. Marine Mammal Science, 21(1), 121–135. Forcada, J., Trathan, P. N., Reid, K., & Murphy, E. J. (2005). The effects of global climate
variability in pup production of antarctic fur seals. Ecology, 86(9), 2408–2417. Friedlaender, A. S., Johnston, D. W., Fink, S. L., & Lavigne, D. M. (2006). Variation in Ice Cover on
the East Coast of Canada , Implications for harp and hooded seals. Environment, 1–8. Friedlaender, A. S., Johnston, D. W., & Halpin, P. N. (2010). Effects of the North Atlantic
Oscillation on sea ice breeding habitats of harp seals (Pagophilus groenlandicus) across the North Atlantic. Progress in Oceanography, 86(1–2), 261–266.
Gilbert, J. R., Waring, G. T., Wynne, K. M., & Guldager, N. (2005). Changes in abundance of
harbor seals in maine, 1981-2001. Marine Mammal Science, 21(3), 519–535. Grémillet, D., Lewis, S., Drapeau, L., Van Der Lingen, C. D., Huggett, J. A., Coetzee, J. C., Verheye,
H. M., Daunt, F., Wanless, S., & Ryan, P. G. (2008). Spatial match-mismatch in the Benguela upwelling zone: Should we expect chlorophyll and sea-surface temperature to predict marine predator distributions? Journal of Applied Ecology, 45(2), 610–621.
Gulland, F. D., & Hall, A. J. (2007). Is marine mammal health deteriorating? Trends in the global
reporting of marine mammal disease. EcoHealth, 4(2), 135–150. Hall, A., & Kershaw, J. (2012). Marine Mammal Scientific Support Review of the status , trends
and potential causes for the decline in abundance of harbour seals around the coast of Scotland, (November).
Halliday, W. D., Insley, S. J., Hilliard, R. C., de Jong, T., & Pine, M. K. (2017). Potential impacts of
shipping noise on marine mammals in the western Canadian Arctic. Marine Pollution Bulletin, 123(1–2), 73–82.
Hamilton, C. D., Lydersen, C., Ims, R. A., & Kovacs, K. M. (2015). Predictions replaced by facts: A
keystone species’ behavioural responses to declining arctic sea-ice. Biology Letters, 11(11), 1–6.
38
Hammill, M. O., Heyer, C. E. den, Bowen, W. D., & Lang, S. C. (2017). Grey Seal Population
Trends in Canadian Waters, 1960-2016 and Harvest Advice. Canadian Science Advisory Secretariat.
Hammill, M. O., Stenson, G. B., Doniol-Valcroze, T., & Mosnier, A. (2015). Conservation of
northwest Atlantic harp seals: Past success, future uncertainty? Biological Conservation, 192, 181–191.
Hanni, K. D., Long, D. J., Jones, R. E., Pyle, P., & Morgan, L. E. (1997). Sightings and Strandings of
Guadalupe Fur Seals in Central and Northern California, 1988-1995. Journal of Mammalogy, 78(2), 684–690.
Harris, D. E., & Gupta, S. (2006). GIS-based Analysis of Ice-breeding Seal Strandings in the Gulf
of Maine. Northeastern Naturalist, 13(3), 403–420. Harris, D. E., Lelli, B., & Jakush, G. (2002). Harp Seal Records From the Southern Gulf of Maine:
1997 – 2001. Northeastern Naturalist, 9(3), 331–340. Harwood, J. (2001). Marine mammals and their environment in the twenty-first century. Journal
of Mammalogy, 82(3), 630–640. Hayes, S. A., Josephson, E., Maze-Foley, K., & Rosel, P. E. (2017). US Atlantic and Gulf of Mexico
Marine Mammal Stock Assessments - 2016. NOAA Technical Memorandum NMFS-NE-241, (June), 274.
Hofman, R. J. (1987). History, goals, and achievements of the regional marine mammal
stranding networks in the United States. Second Marine Mammal Stranding Workshop, 7–16.
Ijsseldijk, L. L., Brownlow, A., Davison, N. J., Deaville, R., Keijl, G., Siebert, U., & Doeschate, M. T.
I. (2018). Spatiotemporal trends in white-beaked dolphin strandings along the North Sea coast from 1991 – 2017. Lutra, 61(1), 153–163.
Johnston, D. W., Bowers, M. T., Friedlaender, A. S., & Lavigne, D. M. (2012). The effects of
climate change on harp seals (Pagophilus Groenlandicus). PLoS ONE, 7(1), 1–8. Johnston, D. W., Frungillo, J., Smith, A., Moore, K., Sharp, B., Schuh, J., & Read, A. J. (2015).
Trends in stranding and by-catch rates of gray and harbor seals along the northeastern coast of the United States: Evidence of divergence in the abundance of two sympatric phocid species? PLoS ONE, 10(7), 1–12.
Katona, S. R., Richardson, D. T., & Rough, V. (1993). A field guide to whales, porpoises, and seals
from Cape Cod to Newfoundland (Fourth Edi). Smithsonian Institution Press.
39
Koschinski, S., Culik, B. M., Henriksen, O. D., Tregenza, N., Ellis, G., Jansen, C., & Käthe, G.
(2003). Behavioural reactions of free-ranging porpoises and seals to the noise of a simulated 2 MW windpower generator. Marine Ecology Progress Series, 265, 263–273. h
Kucklick, J. R., Struntz, W. J., Becker, P. R., York, G. W., O’Hara, T. M., & Bohonowych, J. E.
(1994). Persistent organochlorine pollutants in ringed seals and polar bears collected from northern Alaska. Phytochemical Analysis, 5(5), 261–265.
Laidre, K. L., Stern, H., Kovacs, K. M., Lowry, L., Moore, S. E., Regehr, E. V., Ferguson, S. H., Wiig,
O., Boveng, P., Angliss, R. P., Born, E. W., Litovka, D., Quakenbush, L., Lydersen, C., Vongraven, D., & Ugarte, F. (2015). Arctic marine mammal population status, sea ice habitat loss, and conservation recommendations for the 21st century. Conservation Biology, 29(3), 724–737.
Lavigueur, L., & Hammill, M. O. (1993). Distribution and seasonal movements of grey seals,
Halichoerus grypus, born in the Gulf of St. Lawrence and easter Nova Scotia shore. Canadian Field-Naturalist, 107(3), 329–340.
Lelli, B., Harris, D. E., & Aboueissa, A. M. (2009). Seal Bounties in Maine and Massachusetts,
1888 to 1962. Northeastern Naturalist, 16(2), 239–254. h Li, J., Sun, C., & Jin, F. F. (2013). NAO implicated as a predictor of Northern Hemisphere mean
temperature multidecadal variability. Geophysical Research Letters, 40(20), 5497–5502. Lucas, Z., & Stobo, W. T. (2000). Shark-inflicted mortality on a population of harbour seals
(Phoca vitulina) at Sable Island, Nova Scotia. Journal of Zoology, 252(3), 405–414. Macleod, C. D., Bannon, S. M., Pierce, G. J., Schweder, C., Learmonth, J. A., Herman, J. S., &
Reid, R. J. (2005). Climate change and the cetacean community of north-west Scotland. Biological Conservation, 124, 477–483.
Mannocci, L., Dabin, W., Augeraud-Véron, E., Dupuy, J. F., Barbraud, C., & Ridoux, V. (2012).
Assessing the impact of bycatch on dolphin populations: The case of the common dolphin in the Eastern North Atlantic. PLoS ONE, 7(2), 1–12.
Martínez-Abraín, A. (2008). Statistical significance and biological relevance: A call for a more
cautious interpretation of results in ecology. Acta Oecologica, 34(1), 9–11. Matthiopoulos, J., Smout, S., Winship, A. J., Thompson, D., Boyd, I. L., & Harwood, J. (2008).
Getting beneath the surface of marine mammal-fisheries competition. Mammal Review, 38, 167–188.
40
McAlpine, D. F., Stevick, P. T., Murison, L. D. (1999). Increase in Extralimital Occurrences of Ice-breeding Seals in the Northern Gulf of Maine Region: More Seals or Fewer Fish? Marine Mammal Science, 15(3), 906–911.
Meager, J. J., & Sumpton, W. D. (2016). Bycatch and strandings programs as ecological
indicators for data-limited cetaceans. Ecological Indicators, 60. Moore, M. J., Van Der Hoop, J., Barco, S. G., Costidis, A. M., Gulland, F. M., Jepson, P. D., Moore,
K. T, Raverty, S., & McLellan, W. A. (2013). Criteria and case definitions for serious injury and death of pinnipeds and cetaceans caused by anthropogenic trauma. Diseases of Aquatic Organisms, 103(3), 229–264.
Nakagawa, S., & Cuthill, I. C. (2007). Effect size, confidence interval and statistical significance: A
practical guide for biologists. Biological Reviews, 82(4), 591–605. Olson, D. B. (2002). Biophysical dynamics of ocean fronts. The Sea, 12(January 2002), 187–218. Overholtz, W. J., & Link, J. S. (2007). Consumption impacts by marine mammals, fish, and
seabirds on the Gulf of Maine-Georges Bank Atlantic herring (Clupea harengus) complex during the years 1977-2002. ICES Journal of Marine Science, 64(1), 83–96.
Pace, R. M., Josephson, E., Wood, S. A., Murray, K., & Waring, G. (2019). Trends and Patterns of
Seal Abundance at Haul-out Sites in a Gray Seal Recolonization Zone Trends and Patterns of Seal Abundance at Haul-out Sites in a Gray Seal Recolonization Zone, (March).
Palacios, D. M., Baumgartner, M. F., Laidre, K. L., & Gregr, E. J. (2014). Beyond correlation:
Integrating environmentally and behaviourally mediated processes in models of marine mammal distributions. Endangered Species Research, 22(3), 191–203.
Papastavrou, V., Leaper, R., & Lavigne, D. (2017). Why management decisions involving marine
mammals should include animal welfare. Marine Policy, 79(January), 19–24. Peltier, H., Jepson, P. D., Dabin, W., Deaville, R., Daniel, P., Van Canneyt, O., & Ridoux, V. (2014).
The contribution of stranding data to monitoring and conservation strategies for cetaceans: Developing spatially explicit mortality indicators for common dolphins (Delphinus delphis) in the eastern North-Atlantic. Ecological Indicators, 39, 203–214.
Pershing, A. J., Alexander, M. A., Hernandez, C. M., Kerr, L. A., Bris, A. Le, Mills, K. E., Nye, J. A.,
Record, N. R., Scannell, H. A., Scott, J. D., Sherwood, G. D., & Thomas, A. C. (2016). Response to comments on "Slow adaptation in the face of rapid warming leads to collapse of the Gulf of Maine cod fishery. Science, 352(6284), 423.
41
Pierce, G. J., Santos, M. B., Smeenk, C., Saveliev, A., & Zuur, A. F. (2007). Historical trends in the incidence of strandings of sperm whales (Physeter macrocephalus) on North Sea coasts: An association with positive temperature anomalies. Fisheries Research, 87(2–3), 219–228.
Prado, J. H. F., Mattos, P. H., Silva, K. G., & Secchi, E. R. (2016). Long-term seasonal and
interannual patterns of marine mammal strandings in subtropical western South Atlantic. PLoS ONE, 11(1), 1–23.
Pyenson, N. D. (2011). The high fidelity of the cetacean stranding record: insights into
measuring diversity by integrating taphonomy and macroecology. Proceedings of the Royal Society B: Biological Sciences, 278(1724), 3608–3616.
R Development Core Team 3.0.1. (2013). A Language and Environment for Statistical
Computing. R Foundation for Statistical Computing. Vienna, Austria. Retrieved from http://www.r-project.org
Read, A. J. (2008). The looming crisis: interactions between marine mammals and fisheries.
Journal of Mammalogy, 89(3), 541–548. Reddy, M. L., Dierauf, L. A., & Gulland, F. M. (2001). Marine mammals as sentinels of ocean
health. Marine Mammal Medicine, 3–13. Reijnders, P. H. (1986). Reproductive failure in common seals fedding on fish from polluted
coastal waters. Nature, 324(4), 456–457. Richards, S. A. (2005). Testing ecological theory using the information-theoretic approach:
Examples and cautionary results. Ecology, 86(10), 2805–2814. Roman, J., Altman, I., Dunphy-Daly, M. M., Campbell, C., Jasny, M., & Read, A. J. (2013). The
Marine Mammal Protection Act at 40: Status, recovery, and future of U.S. marine mammals. Annals of the New York Academy of Sciences.
Ruest, B., Neumeier, U., Dumont, D., Bismuth, E., Senneville, S., & Caveen, J. (2015). Recent
wave climate and expected future changes in the seasonally ice-infested waters of the Gulf of St. Lawrence, Canada. Climate Dynamics, 46(1–2), 449–466.
Savenkoff, C., Swain, D. P., Hanson, J. M., Castonguay, M., Hammill, M. O., Bourdages, H.,
Morissette, L., & Chabot, D. (2007). Effects of fishing and predation in a heavily exploited ecosystem: Comparing periods before and after the collapse of groundfish in the southern Gulf of St. Lawrence (Canada). Ecological Modelling, 204(1–2), 115–128.
Schots, P. C., Bue, M. E., & Nordøy, E. S. (2017). Hooded seal (Cystophora cristata) pups ingest
snow and seawater during their post-weaning fast. Journal of Comparative Physiology B: Biochemical, Systemic, and Environmental Physiology, 187(3), 493–502.
42
Sergeant, D. E. (1991). Harp Seals, Man and Ice. Canadian Special Publication of Fisheries and
Aquatic Sciences, 114. Sherman, B. J. (2000). Marine ecosystem health as an expression of morbidity, mortality and
disease events. Seas at the Millennium - an Environmental Evaluation - Volume 3, 41(00), 211–234.
Simeone, C. A., Gulland, F. M. D., Norris, T., & Rowles, T. K. (2015). A systematic review of
changes in marine mammal health in North America, 1972-2012: The need for a novel integrated approach. PLoS ONE.
Simmonds, M. P. (2017). Of Poisons and Plastics: An Overview of the Latest Pollution Issues
Affecting Marine Mammals. In Marine Mammal Welfare (pp. 27–37). Springer. Soulen, B. K., Cammen, K., Schultz, T. F., & Johnston, D. W. (2013). Factors Affecting Harp Seal
(Pagophilus groenlandicus) Strandings in the Northwest Atlantic. PLoS ONE, 8(7). Stevick, P. T., & Fernald, T. W. (1998). Increase in Extralimital Records of Harp Seals in Maine
Northeastern Naturalist, 5(1), 75–82. Swart, R. L., Ross, P. S., Vedder, L. J., Timmerman, H. H., Heisterkamp, S., Loveren, H. V., Vos, J.
G., Reijnders, P. J., & Osterhaus, A. D. (1994). Impairment of Immune Function in Harbor Seals (Phoca vitulina) Feeding on Fish from Polluted Waters. Ambio, 23, 155–159.
Thomas, A. C., Pershing, A. J., Friedland, K. D., Nye, J. A., Mills, K. E., Alexander, M. A., Record, N.
R., Weatherbee, R., & Henderson, M. E. (2017). Seasonal trends and phenology shifts in sea surface temperature on the North American northeastern continental shelf. Elem Sci Anth, 5(2007), 48.
Truchon, M. H., Measures, L., Brêthes, J. C., Albert, É., & Michaud, R. (2018). Influence of
anthropogenic activities on marine mammal strandings in the estuary and northwestern Gulf of St. Lawrence, Quebec, Canada, 1994–2008. Journal of Cetacean Research and Management, 18(October), 11–21.
Truchon, M. H., Measures, L., L’Hérault, V., Brêthes, J. C., Galbraith, P. S., Harvey, M., Lessard,
S., Starr, M., & Lecomte, N. (2013). Marine Mammal Strandings and Environmental Changes: A 15-Year Study in the St. Lawrence Ecosystem. PLoS ONE, 8(3).
Tweedie, M. C. (1984). An index which distinguishes between some important exponential
families. Statistics: Applications and New Directions: Proc. Indian Statistical Institute Golden Jubilee International Conference, 579, 579–604.
43
Vanderlaan, A. S. M., & Taggart, C. T. (2007). Vessel collisions with whales: The probability of lethal injury based on vessel speed. Marine Mammal Science, 23(1), 144–156.
Wares, J. P., Gaines, S. D., & Cunningham, C. W. (2001). A comparative study of asymmetric
gene flow across a marine biogeographic boundary. Evolution, 55(2), 295–306. Waring, G. T., DiGiovanni Jr., R. A., Josephson, E., Wood, S., & Gilbert, J. R. (2015). 2012
Population Estimate for the Harbor Seal ( Phoca vitulina concolor ) in New England Waters, (August).
Williams, R., Gero, S., Bejder, L., Calambokidis, J., Kraus, S. D., Lusseau, D., Read, A. J., &
Robbins, J. (2011). Underestimating the damage: Interpreting cetacean carcass recoveries in the context of the Deepwater Horizon/BP incident. Conservation Letters, 4(3), 228–233.
Wilson, S. C., Trukhanova, I., Dmitrieva, L., Dolgova, E., Crawford, I., Baimukanov, M.,
Baimukanov, T., Ismagambetov, B., Pazylbekov, M., Jüssi, M., & Goodman, S. J. (2017). Assessment of impacts and potential mitigation for icebreaking vessels transiting pupping areas of an ice-breeding seal. Biological Conservation, 214(August), 213–222.
Wood, S. A., Murray, K. T., Josephson, E., & Gilbert, J. (2020). Rates of increase in gray seal (
Halichoerus grypus atlantica ) pupping at recolonized sites in the United States , 1988 – 2019, Journal of Mammalogy, 101(1), 121–128.
Zuur, A. F., Ieno, E. N., & Elphick, C. S. (2010). A protocol for data exploration to avoid common
statistical problems. Methods in Ecology and Evolution, 1(1), 3–14. Zuur, A. F., Ieno, E. N., Walker, N. J., Saveliev, A. A., & Smith, G. M. (2009). Mixed Effects Models
and Extensions in Ecology with R. PhD Proposal (Vol. 1).
44
APPENDIX
Appendix A. Marine mammal stranding response organizations
Organization Address Phone Number College of the Atlantic’s Allied Whale
105 Eden St, Bar Harbor, ME 04609
(207) 288-5644
National Marine Fisheries Service 130 Oak St, Ellsworth, ME 04605
(207) 664-0508
Maine Department of Marine Resources
32 Blossom Ln, Augusta, ME 04330
(207) 624-6550
Marine Mammals of Maine P.O. Box 751, Bath, ME 04530 (207) 844-8718
University of New England Marine Animal Rehabilitation Center*
11 Hills Beach Rd, Biddeford, ME 04005
N/A
Marine Animal Lifeline* New Hampshire N/A Seacoast Science Center 570 Ocean Boulevard
Rye, NH 03870 (603) 997-9448
New England Aquarium 1 Central Wharf, Boston, MA 02110 (617) 973-5200
International Fund for Animal Welfare
290 Summer Street, Yarmouth Port, MA 02675
(202) 536 1900
Riverhead Foundation 467 E Main St, Riverhead, NY 11901
(631) 369-9840
National Aquarium in Baltimore 501 E Pratt St, Baltimore, MD 21202
(410) 576-3880
*No longer in operation
45
BIOGRAPHY OF THE AUTHOR
Holland Haverkamp has a professional background in filmmaking and photography, but
has long been interested, concerned and passionate about the health of our planet’s ecologies,
both marine and terrestrial. He is guided by a notion that all life and non-life (should there be
such a thing) are intertwined, never acting independently. Holland and his partner have six
children, whom create a full and delightfully overwhelming life for them all. He is a candidate
for the Master’s degree in Ecology and Environmental Sciences from the University of Maine in
August, 2020.